Environmental assessment of Mill creek in the vicinity of the Port Elgin landfill site, Bruce County.

BioMAP Report SWR-3

Ministry of Environment and Energy

Southwestern Region

Water Resources Assessment Unit

985 Adelaide St. South

London, Ontario N6E-1V3

ENVIRONMENTAL ASSESSMENT OF MILL CREEK
IN THE VICINITY OF THE PORT ELGIN LANDHLL SITE,

BRUCE COUNTY

J.D. Westwood & Ronald W. Griffiths

c.l
a aa

June 1994

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Table of Contents

Page

Executive Summary ii

Introduction t

Materials and Methods 1

Results 2

Disciission 3

Acknowledgements 5

References 6

Tables 8

Figures 12

BioMAP i Westwood & Griffiths, 1994

EXECUTIVE SUMMARY

The Southwestern Region of the Ministry of Environment and Energy conducted an
environmental assessment in August of 1993 to document the ecosystem health of Mill Creek in the
vicinity of the Port Elgin Landfill Site and determine if leachate from the landfill was affecting
water quality. Toxic conditions were not evident in the stretch of Mill Creek receiving leachate.
The noticeable growth of filamentous green algae, however, suggests that the leachate may have a
localized nutrient enrichment effect on the stream ecosystem. The benthic macroinvertebrate faima
found throughout the study area was indicative of an nutrient -enriched, warm -water stream. The
wide occurrence of agriculture in the drainage basin and storm-water drainage from the Port Elgin
area likely account for the impaired health of the creek.

BioMAP u Westwood & Griffiths, 1994

INTRODUCTION

The Port Elgin Landfill Site is located to the east of Port Elgin, Ontario, adjacent to the
sewage treatment plant and consists of a closed (old) landfill site and an active (new) landfill site
(Figure 1). Dames and Moore, Canada Limited (1993) noted that a plume of leachate containing
chlorides, ammonia and iron was migrating ftx>m the Port Elgin Landfill Site towards Mill Creek,
which flows along the eastern boundary of the landfill site. Because the leachate could enter the
creek through groundwater inputs and disrupt the aquatic community, a concern was raised
regarding the water quality risk from the advancing leachate plume from both the old and new
landfill sites. Ammonia concentrations of up to 13 mg/L were noted from observation wells near
the creek in the late 1980's (Morrison Beatty 1991); ammonia is a major concern because it
suggests anaerobic conditions within the groundwater and is lethally toxic to aquatic life at low
concentrations (Hellawell 1986). In response, the Southwestern Region of the Ministry of
Environment and Energy conducted an envirormiental assessment to document the ecosystem
health of Mill Creek in the vicinity of the landfill site and determine if leachate from the landfill was
affecting water quality.

MATERIALS AND METHODS

To assess the water quality of Mill Creek in the vicinity of the Port Elgin landfill site, three
sampling sites were established along the creek (Figure I). Site 1 was located upstream of the
landfill site and was assumed to represent reference water quality conditions. Site 2 was located in
a stretch of the stream where the leachate plume from the old landfill site was suspected to enter
Mill Creek Site 3 was located downstream of the plumes from the landfill sites and possible
overflows from the sewage treatment plant. Treated sewage from the sewage treatment plant is not
discharged to Mill Creek, but is piped under the creek and discharged to the Saugeen River. No
farther sites were located downstream of Site 3 because of obvious impacts on the stream caused
by cattle with unlimited access.

Samples of benthic tnacroin vertebrates and water were collected between August 16 and
18, 1993. Standard BioMAP sampling procedures were used to sample the benthic fauna
(Griffiths 1993); two quantitative samples, collected with a Surber sampler enclosing a 0.09 m^
area, and a single 30-minute qualitative sample (bucket and sieve) were taken at each site. The

BioMAP 1 Westwood & Griffiths, 1994

Surber sampler had a 600-fi mesh collecting net . The benthos were sorted alive from the debris
and preserved in 80% ethanol. The processed samples were transported to the Southwestern
Regional office in London for identification.

Water samples were collected at each site on August 1 8 and analyzed at the Southwestern
Regional Laboratory in London for: anunonia, total Kjeldahl nitrogen, nitrite, nitrate, total
phosphorus, dissolved reactive phosphorus, pH, conductivity, and chloride.

Observations of stream characteristics, plant and algae growth, fish and wildlife were noted
throughout the study area. Stream characteristics were also recorded using photography and
video. Water temperature and conductivity were measured in the field. A Magellan 5000 GPS unit
was unit to determine the UTM co-ordinates of the sampling sites.

RESULTS

Mill Creek near the landfill site was characterized by even-flow sections dispersed with
riffle areas. The stream width varied between 2.6 and 9.5 m. Water depths ranged from 5 cm in
riffles to 2 m in poob. The bottom of the stream was composed of small boulders, cobble, gravel
and sand. The stream banks exhibited erosional damage; many gravel and sand bars were present
in the floodplain indicating that the stream periodically experienced high flows. These conditions
were most evident at sites 2 and 3. The riparian habitat was generally forested, except for a small
stretch of meadow between sites I and 2.

The water was clear with a temperature of 23° C at all sites. Phosphorus concentrations
were similar among sites, whereas conductivity, nitrate and chloride concentrations increased from
Site 1 to Site 3 (Table 1). In contrast, ammonia concentrations declined from Site I to Site 3.

At Site 1, located upstream of the County Road#17 bridge (Figures 1 & 2), the substrate
was composed of small boulders, cobble, gravel and sand (Figure 3). Sparse moss and diatom
growth covered the cobble. Marl (travertine) was deposited over the larger cobble, likely
associated with the growth of mosses and algae (e.g. diatoms). At Site 2, the substrate was
composed of cobble, gravel and sand (Figure 2). The filamentous green alga, Cladophora,
covered approximately 60% of the riffle area, but the fronds (filament length) were only a few
centimetres long. A beaver was completing a dam approximately 150 m upstream. At Site 3, the

BioMAP 2 Westwood & Griffiths, 1994

substrate was composed of small cobble, gravel and sand (Figure 2). Pronounced iron staining
(orange colour) was noted over portions of the substrate. Riffle areas were about 60% covered
with Cladophora stubble. Spyrogyra was common in even-flow areas, beginning downstream of
Site 2 and continuing downstream of Site 3 (Figure 3),

Macroinvertebrate densities were similar among sites, ranging from 700 to 1200 per 0.09
m^ (Figure 4). Species richness was also similar among sites; the number of taxa per 0.09 m^
(alpha richness) ranged from 30 to 37 (Figure 4) while the number of taxa per site (gamma
richness) ranged from 48 to 54. A total of 80 taxa was collected throughout the study area (Table
2). Insects accounted for 98% of the benthic fauna at sites 1 and 2 and 94% of the fauna at Site 3.
Worms were not found at Site 1, but accounted for 1 % and 4.5% of the fauna at sites 2 and 3,
respectively. Filter-feeding macrojuvertebrates (e.g. Cheumatopsyche, Hydropsyche,
Microtendipes, tanytarsinid midges, clams) increased from 55% of the fauna at Site 1 to 72% of
the fauna at sites 2 and 3, whereas scrapers (e.g. Helicopsyche, heptageniid mayflies, psephenid
beetles, snails) declined from 29% of the fauna at Site 1 to 15% of the fauna at Site 3. A shift in
species composition was also noted: baetid mayflies, Stenonema pulchellum, Stenonema
mediopunctatum , and lumbriculid worms increased in density from Site 1 to Site 3, while
Petrophila, Stenelmis crenata, Psephenus herricld , flatworms, and the dipt erans: Microtendipes,
empidids, tipulids, athericids, declined in density from Site 1 to Site 3 (Table 2).

Fish were present throughout the study area; rock bass (AmblopUtes rupestris), white
sucker (Castostomus commersoni), common shiner (Notropis comutus), creek chub (Semotilus
atromaculatus)^ darters (Etheostoma) and a northern brook lamprey (Ichthyomyzon fossor)
specifically were observed. The green frog (Rana clamitans) and the northern leopard frog (Rana
pipiens) were noted throughout the floodplain. Frogs were also observed in the pond located
between the old landfill site and Mill Creek. The water in the pond had a conductivity of 630 juS
and temperature of 24° C.

DISCUSSION

The higher chloride concentrations at sites 2 and 3 (approximately 14 mg/L) relative to Site
1 (8 mg/L) implies that leachate from the Port Elgin landfill site is gaining access to Mill Creek via
groundwater inflow. Toxic conditions, however, were not evident in tiiis stretch of Mill CreeL
Macroinvertebrate density and species richness at sites 2 and 3 were not less than that found at the

BioMAP 3 Westwood& Griffiths, 1994

reference site (Site 1). In addition, the abundance of species sensitive to metal concentrations,
such as baetid and heptagenid mayflies (Clements 1994; Clements et al. 1992), actually increased
from Site 1 to Site 3. The observed occurrence of frogs and fishes throughout the study area
similarly suggests that the leachate entering the creek was not having toxic effects on the aquatic
biota.

The benthic macroinvertebrate fauna found throughout the study area is indicative of an
nutrient-enriched, warm-water stream. The density of macroinvertebrates in similar sized,
unimpaired (healthy) streams in Grey and Bruce Counties typically range from 100 to 500
organisms per 0.09 m^ (Westwood 1982, 1983; Griffiths, unpubl. data). The macroinvertebrate
density in the study area of Mill Creek was 50% to 1 50% higher than the maximum density noted
in unimpaired streams. The wide occurrence of agricultiire in the drainage basin and storm- water
drainage from the Port Elgin area likely account for the impaired health of the creek.

The noticeable growth of filamentous green algae downstream of Site 2, however, suggests
that the leachate may have a localized nutrient enrichment effect on the stream ecosystem.
Ammonia concentrations ranging up to 13 mg/L have been measured in water samples from
observation wells near the creek during the late 1980's (Morrison Beatty 1991). The average
ammonia concentration in the groundwater near the creek was estimated to be 0.2 mg/L in 1993
(Dames and Moore, Canada Limitedl994), about an order of magnitude greater than that measured
in the creek (Table 1). Similar growth of filamentous green algae has been observed in the
Bighead River adjacent to the Meaford landfill site (Griffiths, personal observation), in the Rocky
Saugeen River adjacent to a landfill site near Markdale (Westwood, personal observation), and in
the Middle Thames River downstream of a rendering facility that infiltrated ammonia-enriched
wastewaters adjacent to the river (Griffiths, personal observation).

The occurrence of filamentous algae at sites 2 and 3 probably accounts for many of the
differences observed in the community structure of the benthic fauna relative to Site 1 .
Filamentous algae is a food resource to some macroinvertebrates, provides food resources in the
form of periphyton, growing on the stands of the filamentous algae, and organic matter filtered
from the stream for others, provides attachment surfaces for filter-feeders, increases habitat
heterogeneity by slowing currents, trapping detritus, blocldng light, altering dissolved oxygen
concentrations and daily pattern, and excludes some taxa by occupying attachment sites (Dudley et
al. 1986). The higher abundance of baetid and heptagenid mayflies and lumbriculid worms at sites
2 and 3 probably reflects the increased availability of periphyton and organic matter provided by

BioMAP 4 Westwood & Griffiths, 1994

tlie filamentous algae and the protection afforded by the algae from strong currents. The reduced
proportion of scrapers noted at sites 2 and 3, particularly Stenelmis, Psephenus herricki,
HeUcopsyche and Petrophila, probably reflects the reduced availability of open space habitat used
by these taxa because of the growth of the algae. The higher proportion of filter-feeding
macroinvertebrates at sites 2 and 3, such as the caddisfiies: Hydropsyche, Chimarra, Psychomyia,
and the midges: tanytarsini, Microtendipes, probably reflects the increased availability of stable
attachment points for their nets provided by the algal mats. The greater proportion of filter- feeders
at sites 2 and 3 is probably a result of the greater availability of seston (food) in the stream
produced in the more lentic waters observed through the "meadow section" of the stream and
behind the beaver dam; the closer proximity of Site 2 to this source of food likely accounts for the
higher density of filter-feeders relative to Site 3. The lower abundance of flatworms at sites 2 and
3 possibly reflects the reduced area of open space habitat and increased siltation which fouls their
mucus-trail traps, reducing their ability to catch prey.

In conclusion, the leacbate currently entering Mill Creek from the Port Elgin Landfill Site is
not toxic to aquatic life. The occurrence of filamentous green algae, however, suggests that the
leachate is likely having a localized nutrient-enrichment effect on the stream ecosystem.
Differences in the benthic macroinvertebrate fauna relative to an upstream reference site appear
largely to be a result of the filamentous algae modifying habitat conditions.

ACKNOWLEDGEMENTS

We gratefully acknowledge the dedicated field work of Mike Johns and Annette Jones. We
also appreciate the comments provided by Denis Veal and Doug Huber on an earlier version of this
paper.

BioMAP 5 Westwood & Griffiths, 1994

REFERENCES

Clements, W.H. 1994. Benthic invertebrate community responses to heavy metals in the Upper
Arkansas River Basin, Colorado. J. N. Am. Benthol. Soc. 13: 30-44.

Clements, W.H., D.S. Cherry, and J.H. van Hassel. 1992. Assessment of the impact of heavy
metab on benthic communities at the Clinch River (Virginia): evaluation of an index of
coimnunity sensitivity. Can. J. Fish. Aquat. Sci. 49: 1686-1694.

Dames and Moore, Canada Limited. 1993. Town of Port Elgin Landfill Site 1992 Monitoring
Report. Prepared for the Town of Port Elgin. Prepared by Dames and Moore Canada
Limited, Mississauga, Ontario.

Dames and Moore, Canada Limited. 1994. Town of Port Elgin Landfill Site 1993 Monitoring
Report. Prepared for the Town of Port Elgin. Prepared by Dames and Moore Canada
Limited, Mississauga, Ontario.

Dudley, T.L., S.D. Cooper, and N. Hemphill. 1986. Effects of macroalgae on a stream
invertebrate conmiunity. J. N. Am. Benthol. Soc. 5: 93-106.

Hellawell, J.M. 1986. Biological indicators of freshwater pollution and envirotunetttal
management. Elsevier Applied Science Publ., New York, N.Y. 546 pp.

Griffiths, R.W. 1993. BioMAP: Concepts, Protocols and Sampling Procedures for the

Southwestern Region of Ontario. BioMAP Report SWR-1. Ministry of Environment and
Energy, Southwestern Region. 30 pp.

Morrison Beatty. 1991. 1990-1991 Monitoring Report for the Town of Port Elgin Landfill Site.
Prepared for the Town of Port Elgin. Prepared by Morrison Beatty (A Division of Trow,
Dames and Moore), Mississauga, Ontario,

Westwood, J.D. 1982. Water quality and hydrology of the Bighead River, Grey County. Ministry
of the Environment, Southwestern Region. London, Ontario.

BioMAP 6 Westwood & Griffiths, 1994

Westwood, J.D. 1983. Water quality and hydrology of the Beaver River, Grey County. Ministry
of the Environment, Southwestern Region. Lx)ndon, Ontario.

BioMAP 7 Westwood & Griffiths, 1994

Table 1: Water chemical characteristics at 3 sites along Mill Creek. Water samples
were collected on August 18, 1993. See Figure 1 for locations of sites.

Chemical Variables

SITE1

SITE 2

SITE 3

Location (UTM)

4 919 677 N

4 920 344 N

4 920 520 N

469 820 E

470 674 E

470 830 E

Ammonia-N (mg/L)

0.041

0.030

0.026

Total Kjeldahl Nitrogen (mg/L)

0.56

0.44

0.47

Nitrite-N (mg/L)

0.01

0.02

0.02

Nitrate-N (mg/L)

0.9

1.1

1.5

Total Phosphorus (mg/L)

0.016

0.017

0.012

Dissolved Reactive Phosphorus (mg/L)

<0.001

<0.001

<0.001

pH

7.98

7.88

7.93

Conductivity (|uS)

521

559

561

Chloride (mg/L)

8.0

14.1

13.7

BioMAP

8

Westwood & Griffiths, 1994

Table 2: Mean density of benthic macroinvertebrates (number per 09 sq. m) at 3 sites
along Mill Creek collected from August 16-18, 1993 P denotes that the taxon
was present at the site. See Figure 1 for location of sites.

Sites
12 3

Insects:
ALDERFLIES:
Siaiidae:
Sialis
AQUATIC MOTHS:
Lepidoptera
Pyralidae:
Petrophila

62

BEETLES:
Dytiscidae:

Deronectes

Hydroporus
Elmidae:

Dubiraphia bivittata

Oubiraphia vittata

Macronychus glabratus

Microcylloepus pusillus

Optioservis

Optioservis fastiditus

Optioservis trivittatus

Stenelmis

Stenelmis crenata
Haliplidae:

Peltodytes
Hydrophilidae:

Berosus

Heiopliorus
Psephenidae:

Ectopria

Psephenus herricki
BUGS:
Corixidae:

Sigara
Gerridae:

Limnoporus
CADDISFLIES:
Helicopsychidae:

Helicopsyche
Hydropsychidae:

Cheumatopsyche

Hydropsyche
Hydroptilidae;

Hydroptila
Leptocetidae:

Oecetis
Umnephilidae:

Hydatophylax

Neophylax

Pycnopsyche

:lV^«^^»5;»«lt'4'*W«M-,^» +i''*^W- < \< V*> ^ '

P

6.5
0.5

7

1.5

0.5

138.5

6

0.5
47

13.5

0.5

P

6

0.5

22.5
3.5
12.5
23
2.5

0.5

0.5

0.5

6

8.5
P

0.5
24

2

11.5

1.5

P
1

0.5

P

P

32

119.5

6

288
71.5

329
385.5

338
60

1

2

1

1.5

2

1

P

P

P

BioMAP

Westwood & Gnffiths, 1994

Table 2: continued.

Sttes
2

Philopotamidae:
Chimarra 62 102 54

Polycentropodidae:
Neureclipsis 1

Polycentropus P

Psychomyiidae:
Psychomyia 5 1

DAMSELFLIES;

Calopterygidae;
Calopteryx maculata

Coenagrionidae
DRAGONFLIES:

Aeshnidae:

Basiaeschna P

Boyeria P

MAYFLIES;

Baetidae:

Acentrella ample 2 6.5

Acerpenna pygmaeus 11 6.5 13.5

Baetissp.C P 9.5 20.5

Baetis spp. 2 2.5 18

Centroptilum (ss) P P

Caenidae:
Caenis 0.5 6.5 0.5

Ephermerellidae:
Seratella 4.5

Ephemeridae:
Ephemera simulans P

Heptageniidae:
Stenacron interpunclatum 1.5 P 0.5

Stenonema femoratum P P

Stenonema mediopunctatum P 0.5 15

Stenonema pulchellum P 2.5

Stenonema sp.A 0.5

Stenonema 1 1-5 6.5

Oligoneuriidae:
Isonychia 4.5 1.5

Tricoryttiidae:
Tricxjrythodes 0.5

TRUE FLIES; (^

Athencidae;
Atherix 1.5 0.5

Chironomidae:

Chironomini 26.5 38 21

ChironominJ Genus A 1

Cryptochironomus 1 1

Microtendipes 44.5 35.5 4.5

Tanytarsini 15 34 16

Orthocladiinae 4.5 7 13

Pentaneurini 20.5 20.5 9

Monodiamesa 0.5

BioMAP 10 Westwood& Griffiths, 1994

Sites

1

2

3

4

2.5

0.5
0.5

1

0.5
1

2

0.5

Table 2: continued.

Empididae:

Hemerodromia
Simuliidae
Tipulidae:

Antocha

Hexatoma

Tipula

Crustaceans:

AMPHIPODS: J^

Gammaridae:
Gammarus 0.5 1

Talitndae:

Hyalella azteca 0.5 2

CRAYRSHES:
Astacidae:

Orconectes propinquus P P P

ISOPODS:
Asellidae:
Caeddotea 0.5

Molluscans:

Sphaenidae:

Sphaerium 6.5 1 0.5

SNAILS:
Ancylidae:

Ferrissia 0.5 1 5

Hydrobiidae:

Amnicxila P P

Physidae:

Physella 1 1 P

Planorbidae:

Gyraulus P

Helisoma anceps P

Valvalidae:

Valvala tricarinata P P

Annelids:

WORMS: sMi^'^^is^^ilisd^^

Lumbriculidae 18 32

LEECHES:

Glossiphonidae:
Placobdella parasitica P

Phylum Platyheiminthes:
iPATWORMS:
Tridadida 9.5 2.5

Organisms per Sample 883 1236 708

Taxa per Sample 30.5 36.5 33.5

Taxa per Site 48 51 54

BioMAP 11 Westwood & Gnffiths, 1994

250 500 750 1000 m

Figure 1: Location of the biological sampling sites along Mill Creek, August 1993.

BioMAP

12

Westwood & Griffiths, 1994

Figure 2: Pictures of sampling sites 1 , 2, and 3 along Mill Creek.

BioMAP

13

Westwood & Griffiths, 1994

Figure 3: Pictures of the stream bottom at Site 1 (upper) and filamentous algae
between sites 2 and 3 along Mil! Creel<.

BioMAP

14

Westwood & Griffiths. 1994

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Figure 4: Species richness (upper graph) and macroinvertebrate density (lower
graph) at 3 sampling sites along Mill Creek, August 1993, Error bars represent
1S.D. See Figure 1 for location of sampling sites.

BioNfAP

15

Westwood & Griffiths, 1994

BioMAP Reports available from
the Ministry of the Environment and Energy, Southwestern Region, London, Ontario.

1. Program Reports:

Griffiths, RW. 1993. BioMAP: Concepts, Protocols and Sampling Procedures for the
Southwestern Region of Ontario. BioMAP Report SWR-1. 30 pp.

2. Water Quality Assessment Reports:

Westwood, J.D. and M. Johns. 1993. Environmental Assessment of the Teeswater River at the
VillageofTeeswater, Bruce County. BioMAP Report SWR-2. 22 pp.

Westwood, J.D. and R.W. Griffiths. 1994. Environmental Assessment of Mill Creek in the

vicinity of the Port Elgin Landfill Site, Bruce Coimty. BioMAP Report SWR-3. 15 pp.

(7393)
MOE/ENV/AITB

Date Due

MOE/ENV/AITB
Westwood, J.
Environmental
of Mill creek
c.

assessment
in the aitb
1 a aa